Birds are commonly used as an example of the strongly declining farmland biodiversity in Europe. The populations of many species have been shown to suffer from intensification of management, reduction of landscape heterogeneity, and habitat loss and fragmentation. These conditions particularly dominate farmland in the economically well developed countries of Western Europe. Currently, the farmland environment in Central-Eastern Europe is generally more extensive than in Western Europe and a larger proportion of people still live in rural areas; thus generating different conditions for birds living in agricultural areas. Furthermore, the quasi-subsistence farming in much of Central-Eastern Europe has resulted in agricultural landscapes that are generally more complex than those in Western Europe. To protect declining bird populations living in farmland, detailed knowledge on both species and communities is necessary. However, due to scientific tradition and availability of funding, the majority of studies have been carried out in Western Europe. In consequence this provokes a question: are findings obtained in western conditions useful to identify the fate of farmland bird biodiversity in Central-Eastern Europe? Therefore, the major goal of this paper is to highlight some local and regional differences in biodiversity patterns within EU farmland by comparing intensive agricultural landscapes with more extensive ones. More specifically, we aim to outline differences in agricultural landscapes and land use history in the two regions, use farmland birds to provide examples of the differences in species dynamics and species-habitat interactions between the two regions, and discuss possible social and ecological drivers of the differences in the context of biodiversity conservation. Factors governing spatio-temporal dynamics of farmland bird populations may differ in intensive and extensive landscapes as illustrated here using the Grey Partridge Perdix perdix and the Red-backed Shrike Lanius collurio as examples. The unevenness of farmland bird studies distribution across Europe was also presented. We call for more emphasis on pluralism in furthering both pan-European research on farmland bird ecology and conservation strategies. We also highlight some features specific to Central-Eastern Europe that merit consideration for the more efficient conservation of farmland birds and farmland biodiversity across Europe.
FARMLAND BIODIVERSITY AND ITS CONSERVATION WITHIN THE EUROPEAN UNION
Farmland biodiversity is currently under threat in much of Europe. Declines in both species numbers and in population sizes have been recorded in all major taxa including plants (e.g. Andreasen et al. 1996), insects (e.g. Kuussaari et al. 2007, Van Dyck et al. 2009), birds (e.g. Wretenberg et al. 2007), and mammals (de Heer et al. 2005). Some of the major drivers of biodiversity loss in farmland are linked to management intensification (e.g. Tscharntke et al. 2005, Báldi & Faragó 2007) and landuse change (e.g. Orłowski 2004, 2005, 2010, Kuemmerle et al. 2008, Spitzer et al. 2009). The major policy tools available for halting biodiversity loss in farmland are agri-environment schemes and the declaration of protected areas. Although both approaches may be powerful tools for biological conservation in farmland, recent findings showed mixed benefits of agrienvironment schemes for biodiversity. Specifically, they have been demonstrated to be less effective in landscapes highly affected by intensive management (Kleijn et al. 2006, Konvička et al. 2008, Ohl et al. 2008) then in less impacted landscapes (Kovács-Hostyýnszki et al. 2011) and have limited efficiency in promoting small-scale, quasi-subsistence, and often traditional farming. However, the meta-analysis by Batáry et al. (2011) suggested that agri-environment schemes could benefit biodiversity, for example, in simple arable landscapes. The establishment of protected areas (such as the Natura 2000 sites in the EU) may, in turn, result in conflicts with local communities and are therefore suboptimal for management for biodiversity (Kluvánková-Oravská et al. 2009). Moreover, in some Eastern European countries a considerable farmland biodiversity is found outside Natura 2000 areas. For example, the traditional model of field division by perennial field margins, retained in many regions of Poland, significantly improves the biodiversity, irrespective of the protection system (Wuczyński et al. 2011). Recently this value has been threatened, for example by urbanisation, infrastructure development, and the adoption of the Common Agricultural Policy.
Biological conservation in Europe's farmland remains, therefore, a challenge for both conservation biologists and policy makers. To develop truly efficient and large-scale (e.g. the EU or all of Europe) conservation strategies, both researchers and policy makers need to understand regional differences in social and ecological systems and how these are linked to biodiversity.
The major goal of this paper is to highlight some local and regional differences in biodiversity patterns within EU farmland by comparing intensive agricultural landscapes with more extensive ones. More specifically, we aim to (i) outline differences in agricultural landscapes and landuse history in the two regions, (ii) use farmland birds to provide examples of the differences in species dynamics and species-habitat interactions between the two regions, and (iii) discuss possible social and ecological drivers of the differences in the context of biodiversity conservation. In the following, we “divide” Europe into two main regions that differ with respect to the agricultural impact on habitats and landscapes: the EU15 located mainly in Western Europe (Austria, Belgium, Danmark, Finland, France, Germany, Greece, Ireland, Italy, Luxembourg, Portugal, Spain, Sweden, the UK, The Netherlands) and the new member states that joined the EU in 2004 and 2007 and which are located mainly in Central and Eastern Europe (Bulgaria, Cyprus, Czech Republic, Estonia, Hungary, Latvia, Lithuania, Malta, Poland, Romania, Slovakia, Slovenia). Hereafter, we refer to the two regions as “Western Europe” (WE) and “Central-Eastern Europe” (CEE).
Bird communities are regarded as an important group for assessing the extent of land use change on overall biodiversity because they are: (i) flagship species, that are popular with the public and visible on a political arena, (ii) they are relatively easy to survey, and finally (iii) they are sensitive to environmental change, including agricultural intensification (Gregory et al. 2005, 2007, Reif et al. 2008, Sanderson et al. 2009).
AGRICULTURAL LANDSCAPES AND FARMLAND BIRD POPULATIONS IN WESTERN AND CENTRAL-EASTERN EUROPE
Agriculture differs between WE and CEE in terms of its role in society and level of intensification (Table 1). In general, in CEE national agricultural production plays a much more important role in economy and society compared to WE. The proportion of the human population employed in agriculture is several times larger in CEE compared to WE (Table 2). At the same time, CEE countries differ in the outcomes of past agricultural intensification: in some states, such as the Czech Republic and much of Slovakia, the communist “collectivist” agriculture created large monoculture fields, not unlike those in Northwestern Europe (Reif et al. 2008). In many CEE countries though, small family farms have retained smaller field sizes and farming methods remain as they were decades ago. In Poland, nearly half of the > 2.5 million farms are still smaller than 2 ha, and this field mosaic is enriched by a dense network of seminatural field margins (Wuczyński et al. 2011). In some others, such as Hungary or Romania, mixed systems with intensive agriculture exist side-by-side with traditional farming in remote areas. Generally, small farms (< 5 ha) are much more abundant in CEE than in WE, for example, there are over 50 times more such farms in Romania than in the UK and nearly 20 times more in Poland than in Germany (Table 2). Productivity also shows great differences between EU regions. For example, milk yield per cow shows nearly a 3-fold difference and potato yields over a 4-fold difference between CEE and WE countries (Central Statistical Office 2009).
Changed demographic conditions and profitability of agriculture in the CEE countries increased land abandonment. But the rural socioecological systems in CEE countries may still represent important reference points for WE conservation targets (de Heer et al. 2005). For example, many traditional rural communities in CEE still use agricultural techniques little changed in centuries. In such conditions, populations of many endangered birds may be stable and widespread. Such systems require mostly maintenance rather than restoration activities, the latter being more typical of the “Western” type of conservation approach (de Heer et al. 2005, Nagy et al. 2009).
Broad comparison of some characteristic features of extensively (Central and Eastern European — CEE) and intensively managed farmland (Western European — WE). Compiled from various available published data.
However, many CEE countries attempt to copy the WE style of intensive farming regardless of its environmental consequences. The existence of agri-environment schemes (AES) has a relatively minor influence on agricultural development (Nagy et al. 2009). The administrative bureaucracy for payments is too complex for small family farms, thus benefits accrue to large farming companies that tend to be much more intensive.
PATTERNS IN BIRD POPULATION SIZES
Bird species composition and abundance in agricultural landscapes show a distinct pattern along the East-West gradient. Several species inhabiting extensive farmland in Europe, including Species of European Conservation Concern (SPEC), are still much more common in CEE than WE (e.g. Moga et al. 2010). This is also true for the majority of birds included in the Farmland Bird Index (FBI) (Gregory et al. 2005). For instance, BirdLife International (2004) estimates abundance of the Corncrake Crex crex as on 551–559 singing males in France and 2000–3100 in Germany. In comparison, the number of singing males estimated for Poland is 30,000–5,000 and for Romania 44,000– 60,000, both countries being smaller than France and Germany. Furthermore, the abundance of White Stork Ciconia ciconia is estimated as 646– 655 pairs in France and 44,000–46,000 pairs in Poland (although only 4,000–5,000 pairs in Romania) and the Corn Bunting Emberiza calandra is estimated as 8,500–12,200 pairs in the UK and 165,000–225,000 pairs in the similarly-sized Hungary.
Selected characteristics of agriculture in some European countries in 2007 presented for CEE and WE groups in alphabetical order (Central Statistical Office 2009).
However, in some CEE countries, little is known how the ultimate factors linked to habitat intensification drive population declines in different bird species (Stoate et al. 2009).
DIFFERENCES IN BIRD POPULATION DYNAMICS
Similarly, long-term trends in the populations of several farmland bird species differ greatly between WE and CEE (Voříšek et al. 2007, European Bird Census Council, www.ebcc.info). The different levels of habitat and landscape structure caused by agricultural management may mean that both spatial and population ecology models fitted to data collected in WE may be of restricted value in CEE. Further increases in agricultural intensification may affect birds in different, and even contrasting, ways in intensively versus extensively managed landscapes. Moreover, all else (e.g. landscape structure, landuse type) being equal, the temporal exposure to intensive land management may also create different patterns of biodiversity.
Differences in the structure and use of agricultural landscapes between WE and CEE are mirrored in changes in bird population abundance. Here we highlight such contrasts using Grey Partridge Perdix perdix and Redbacked Shrike Lanius collurio populations as an example.
Example 1: Grey Partridge survival. In the UK, agricultural intensification, in particular the intensive use of pesticides, was the primary reason for the decline of this species in the post-war period. The result was an associated decrease in chick survival rate to 20%, and increases in nest predation and the physical destruction of nesting habitats in field margins also contributed (Potts 1980, 1986, Potts & Aebischer 1995). Some declines in chick survival rate were found in Western Poland between the 1960s and 1980s (Panek 1991). However, during 1991–2003 the mean chick survival rate in Poland was still 43% (Panek 2005). A decrease in chick survival rate was recently noted in Poland, but was much smaller than that in the UK. Further studies suggested that an increase of adult (female) and brood losses, caused by increased Red Fox Vulpes vulpes predation, were the primary reasons for a considerable population decline of Grey Partridge in Poland. Changes in nest site availability are believed to be an unimportant factor (Panek 2002, 2005).
The importance of weather conditions in determining short-term population fluctuations in Grey Partridge may be also be different in WE (e.g. the UK: Potts 1986, Potts & Aebischer 1995) and CEE countries (e.g. Poland and Czech Republic: Chlewski & Panek 1988, Panek 1992, Salek et al. 2004). This can be related to the more continental situation of CEE countries. In both countries the mortality of chicks is strongly affected by weather conditions. However, in Poland weather strongly influences winter survival: in extreme winters (e.g. high snow cover, low temperatures) the losses of partridge population can be up to 80–90%, making this species more vulnerable to random weather phenomenon in Central Europe than in the UK (see also Salek et al. 2004).
The above example suggests that the factors underlying population fluctuations may show marked regional differences. Whereas in intensively used farmland (e.g. the UK), population decline can be more related to human activity (land use), in CEE the causes of temporal population fluctuations are currently more complex, and human activity is only one of the drivers and may only indirectly affect the bird populations (e.g., through changing predation levels).
Example 2: Red-backed Shrike site fidelity. Differences between farmland landscape structure in WE and CEE may explain spatial dynamics of farmland bird populations. In the intensive agricultural landscapes of WE, the Red-backed Shrike has a high site fidelity (Jakober & Stauber 1987, Massa & Bottoni 1993, Van Nieuwenhuyse 2000) possibly due to the patchy, isolated character of the breeding habitats which “force” shrikes not to venture into an inhospitable matrix. However, in Polish landscapes the site fidelity of this bird was found to be low and there was a pronounced dynamic in its spatial occurrence. The possible explanation of this finding is the widespread availability of breeding sites (Tryjanowski et al. 2007). In such landscapes, population-related phenomena (e.g., local demographic conditions, food resource use) and other biotic relationships (e.g., predation) may be at least as important as habitat availability in determining spatial patterns of bird occurrence.
THE COMPLEX EFFECTS OF AGRICULTURAL INTENSIFICATION AND LAND ABANDONMENT IN CENTRAL-EASTERN EUROPE
Two contrasting patterns of landuse can be observed in the new EU member states since the collapse of socialism in the 1990s: a further increase in agricultural intensification and land abandonment (Brouwer et al. 1991, Jansen & Hetsen 1991, Deffontaines et al. 1995, Stoate et al. 2009). These have contrasting effects on farmland birds with the harmful effect of intensification being generally more obvious (Tucker & Evans 1997, Tworek 2010). Land abandonment temporarily increases biodiversity of bird populations as fallow land undergoes natural succession (e.g. toward grassland and/or scrub encroachment) and attracts many species (Bignal 1998, Orlowski 2004, 2006, Grzybek et al. 2008, Nagy et al. 2009). Land abandonment also increases landscape heterogeneity e.g. by increase of transitional elements between grasslands and forests, such as shrubs and young trees, and by creating a novel and usually diverse field type in the open landscape (Herzon et al. 2006). In Slovakia this had a highly positive effect on the endangered Lesser Grey Shrike Lanius minor (Krištín et al. 2000). This species benefited from the increased shrub cover and abandoned arable land in a predominantly agricultural matrix that dominated breeding territories. The high arthropod (i.e. food) availability was one key element which attracted the Lesser Grey Shrike to these areas. On the other hand, prey availability was negatively associated with the height and density of plant cover (Schifferli 2001, Romanowski & Zmihorski 2008, Hoste-Danyłow et al. 2010), therefore optimal values of vegetation density will differ according to the taxa and species, and a variation of management regimes may be needed.
The potential positive effects of agricultural land abandonment on biodiversity are obscured by two phenomena: invasion of alien plants and increase of predation. In temperate regions, arable land abandonment results in grassland and eventually, in forests. Once invasive species colonize abandoned land the above mentioned succession process may never occur (Skórka et al. 2007). Some species such as alien Goldenrods Solidago spp. or Reed Phragmites australis negatively influence arthropod population sizes (Skórka et al. 2007, Moron et al. 2009) thus potentially reducing food supplies for birds. Indeed, in a study of birds occurring on abandoned grassland in Poland, Skórka et al. (2010) found that invasion of Goldenrods significantly reduced the number of bird species and their abundance (e.g. Corncrake, Lapwing Vanellus vanellus, Yellow Wagtail Motacilla flava and Skylark Alauda arvensis). A substantial positive effect of the invasion was found for only three species: Whinchat Saxicola rubetra, Marsh Warbler Acrocephalus palustris and the introduced Pheasant Phasianus colchicus (Skórka et al. 2010). More studies on the impact of other invasive species on abandoned semi-natural grassland is urgently needed.
Land abandonment may also attract key predators such as the Red Fox and Magpie Pica pica (Skorka et al. unpublished data). These predators were more common in landscapes with a high share (about 20%) of fallow, resulting in lower survival of artificial nests than landscapes where management practices were present (Skorka et al. unpublished data, Tryjanowski et al. 2002, Ejsmond 2008; but see Kujawa & Łcki 2008). The above examples show that the effects of land abandonment on birds are complex and may be both positive and negative, and the net result will depend on the share of abandoned areas at the landscape scale, and on prior land use. Loss of native grassland may be detrimental to biodiversity (Skórka et al. 2010) while abandonment of arable fields may be beneficial to a range of birds associated with meadows (e.g. Whinchat, Corncrake) and shrubs (e.g. Common Whitethroat Sylvia communis and Red-backed Shrike), and wet habitats (Reed Bunting Emberiza schoeniclus, Marsh Warbler and Common Grasshopper Warbler Locustella naevia (Dombrowski & Golawski 2002, Orlowski 2004, 2005, 2010, Berg & Gustafson 2007, Tryjanowski et al. 2009).
No respective phenomenon has been published for WE. It is plausible that most remaining biologically valuable grassland is managed and that invasive species are therefore kept under better control than in CEE.
SPATIAL DISTRIBUTION OF FARMLAND BIRD STUDIES ACROSS EUROPE
The above requires, among others, a greatly increased research effort in the CEE region so that the regional variation in patterns of biodiversity and driving forces behind population changes can be elucidated and taken into account. Studies dealing with the ecology of farmland birds are unevenly distributed across Europe. A good example is an examination of the publications database “Web of Science” which shows that CEE countries are poorly represented (an exception being Poland), compared to WE, in the literature on farmland biodiversity (Fig. 1). Despite relatively large number of papers addressing links between farmland and birds in Europe the scientific effort is highly diversified among particular countries (Fig. 1). The difference between WE and CEE countries is apparent here. In contrast, the proportion of “farmland papers” among all ornithological papers found in Web of Science for a given country is rather stable and does not show any east-west gradient. Finally, the number of ornithological papers covering farmland is seriously diversified in relation to the number of active farmers in a given country. In WE the number of farmers is lower, whereas the number of papers is much higher than in CEE (Fig. 1).
ARE CENTRAL-EASTERN EUROPE COUNTRIES DESTINED TO FOLLOW THE WESTERN EUROPE PATTERN OF FARMLAND BIODIVERSITY DECLINE?
After the Second World War most of the indices of agricultural production were considerably lower in the CEE countries than in WE (reviewed in Bański 2008; see also Donald et al. 2006). This difference was also present after the fall of socialism and communism, i.e. from the 1990s, when agricultural production started to increase from relatively low levels. For example, in Poland the main indices of agricultural production have risen sharply over the last 20 years, although they still do not match the level observed in the old EU member states (FAOSTAT 2007, Bański 2008; see Table 2). Agricultural intensification caused widespread biodiversity decline in the post-war period in WE countries (Robinson & Sutherland 2002, Benton et al. 2003). The economic and technological isolation of CEE countries during the post-war years might have reduced the rate of decline in farmland biodiversity. However, the situation changed following EU accession. The recent data on bird populations in this region suggests a progressive loss of some species, mainly the open farmland specialists, e.g. Lapwing, Skylark and Grey Partridge (Donald et al. 2006, Goławski 2006, Chylarecki & Jawińska 2007, Voříšek et al. 2007, Orlowski & Ławniczak 2009). A time lag in the agricultural intensification in this part of Europe may therefore mean a repeat of the loss of biodiversity experienced in the older EU countries. This scenario can only be avoided if and when efficient policy tools are in place to counteract the impact of intensification. Funding available for agri-environmental management, requirements to strengthen cross-compliance, and enhanced conservation policy may all contribute to a different trajectory for biodiversity in CEE.
The EU has so far failed to stop biodiversity loss in farmland (Balmford et al. 2005, Pedroli et al. 2007). One reason for this may be in the use of wrongly established reference points by conservation biologists.
The available evidence, modest as it is, suggests that the management solutions developed mainly in WE should not be used as a blanket prescription for the whole of Europe. The concept and approaches of conservation in farmland should be better adjusted to regional patterns and peculiarities. In CEE this includes the high level of biodiversity, widespread occurrence of many species which have fragmented populations in WE, the existence of a “soft matrix” (i.e., extensively managed agricultural landscapes), and the predominance of traditional, farming communities. We stress the need for studies to better understand the ecology of farmland birds in CEE countries and their various links to land use. A great advantage could come, for example, from large pan-European research programmes focusing on population dynamics across the continent but with under-lying regional specificity (positive examples are Greenveins, Agripopes, and EASY EU projects). This could help in designing appropriate conservation actions applicable across Europe with modifications for individual regions, where necessary. Actions and programs aimed to halt biodiversity loss in EU farmlands should not be separated from other political decisions, such as social policy for the human rural population.
This opinion paper was initiated by a round-table meeting of Polish researchers held in Turew in March 2010. We would like to thank Jerzy Karg and the technical team of the Field Station, Institute of Agricultural and Forest Environment PAS for their hospitality. András Baldi was supported by OTKA 81971. Martin Hromada was supported by the grants MSM 6007665801 and OPVaV ITMS26220120023. Tibor Hartel was supported by the Strategic grant POSDRU/89/1.5/S/58852, Project “Postdoctoral programme for training scientific researchers” co-financed by the European Social Fund within the Sectorial Operational Program Human Resources Development 2007– 2013.
Appendix. Authors' contact information:
Institute of Ecology and Botany of the Hungarian Academy of Sciences, Alkotmány út 2–4, Vácrátót, H-2163 HUNGARY, e-mail: email@example.com
Department of Zoology, University of Natural Sciences and Humanities in Siedlce, Prusa 12, 08-110 Siedlce, POLAND, email: firstname.lastname@example.org
Mihai Eminescu Trust, Cojocarilor Str. 10, 545400 Sighisoara, ROMANIA, e-mail: email@example.com
Department of Agricultural Sciences, University of Helsinki, P. O. Box 27, FIN-00014, FINLAND, e-mail: firstname.lastname@example.org
University of South Bohemia, Faculty of Biological Sciences, Branišovská 31, 370 05 České Budëjovice, CZECH REPUBLIC; Department of Ecology, Faculty of Humanities and Natural Sciences & Centre of Excellence for Animal and Human Ecology, University in Prešov, 17th November 1, 081 16 Prešov, SLOVAKIA, e-mail: email@example.com
Faculty of Biological Sciences, University of Zielona Góra, Prof. Z. Szafrana Street 1, 65-561 Zielona Góra, POLAND, e-mail: firstname.lastname@example.org
Institute of Entomology, Czech Academy of Sciences, Branišovska 31, 370 05 České Budejovice, CZECH REPUBLIC; University of South Bohemia, Faculty of Biological Sciences, Branišovská 31, 370 05 České Budějovice, CZECH REPUBLIC, e-mail: email@example.com
Institute of Agricultural and Forest Environment, Polish Academy of Sciences, Bukowska 19, 60-809 Poznań, POLAND, e-mail: firstname.lastname@example.org
Institute of Environmental Sciences, Jagiellonian University, Gronostajowa 7, 30-387 Kraków, POLAND, e-mail: email@example.com
Institute of Agricultural and Forest Environment, Polish Academy of Sciences, Bukowska 19, 60-809 Poznań, POLAND, firstname.lastname@example.org
Polish Hunting Association, Research Station, Sokolnicza 12, 64-020 Czempiń, POLAND, e-mail: email@example.com
Institute of Zoology, Poznán University of Life Sciences, Wojska Polskiego 71 C, 60-625 Poznań, POLAND; Institute of Environmental Sciences, Jagiellonian University, Gronostajowa 7, 30-387 Kraków, POLAND, e-mail: firstname.lastname@example.org
Tim H. SPARKS
Institute of Zoology, Poznań University of Life Sciences, Wojska Polskiego 71 C, 60-625 Poznań, POLAND, e-mail: email@example.com
Department of Behavioural Ecology, Adam Mickiewicz University, Umultowska 89, 61-614 Poznań, POLAND, e-mail: firstname.lastname@example.org
Institute of Zoology, Poznań University of Life Sciences, Wojska Polskiego 71 C, 60-625 Poznań, POLAND, e-mail: email@example.com
Institute of Zoology, Poznań University of Life Sciences, Wojska Polskiego 71 C, 60-625 Poznań, POLAND, e-mail: firstname.lastname@example.org
Institute of Nature Conservation, Polish Academy of Sciences, Mickiewicza 33, 31-120 Kraków, POLAND, e-mail: email@example.com
Institute of Nature Conservation, Polish Academy of Sciences, Lower-Silesian Field Station, Podwale 75, 50–449 Wrocław, POLAND, e-mail: firstname.lastname@example.org
Museum and Institute of Zoology, Polish Academy of Sciences, Wilcza 64, 00-679 Warszawa, POLAND, e-mail: email@example.com